Báo cáo khoa học nông nghiệp " Nutrient recovery by rice crops as a treatment for aquaculture solid waste: crop yield, nutrient status and nutrient budgets " doc

Final Nutrient recovery by rice crops as a treatment for aquaculture solid waste: crop yield, nutrient status and nutrient budgets Cao van Phung 1 1. Cuu Long Rice Research Institute, O’Mon, Cantho Province, Vietnam. Email: caovanphung@hcm.vnn.vn , Nguyen be Phuc 2 , Tran kim Hoang 2 and Bell R.W. 3 2. An Giang University, Long Xuyen, An Giang Province, Vietnam 3. School of Environmental Science, Murdoch University, Murdoch 6150, Australia. Abstract Waste from intensive catfish aquaculture production has become a pollutant of surface waters in the Mekong Delta, Vietnam. In the present study, the aim was to treat the solid waste from catfish ponds in the Mekong Delta by land application to padi fields so that the nutrients could be recovered by rice crops as a fertilizer substitute. A field experiment was commenced in the wet season 2007and continued for 6 consecutive rice crops using three doses of solid wastes (1, 2 and 3 tonne/ha) in combination with 1/3 or 2/3 of the recommended inorganic fertiliser rate (60N-17P-24K in wet season and 80N-17.4P- 49.8K/ha in the dry season in kg/ha). Rice yields were generally similar in all treatments in each of the 6 consecutive crops, except that wet season yields declined by ?? with 1/3 rd the fertiliser dose with only 1 t of solid waste. Moreover, with 3 t of solid waste ha, 1/3 rd fertiliser dose gave higher yields in the dry season than with 2/3 rd dose. With straw removal, generally N and K balances were positive in the wet season when yields were low, but negative in the dry season. With straw retention, all K balances were strongly positive but N balances were only positive with the higher solid waste and N fertiliser rates. Phosphorus balances were always strongly positive. Mean levels of organic C, N, available P, K and Zn increased in soils over the course of 6 rice crops. These results suggest that the fishpond solid waste replaced 1/3 to 2/3 of the fertiliser normally applied 1 Corresponding author Cuu Long Rice Research Institute, O’Mon district, Cantho city-Vietnam. Phone No (84) 710861452. Fax: (84) 710861457. Email: caovanphung@hcm.vnn.vn and confirmed that solid wastes from fishponds can be recycled for rice culture to mitigate pollution of waterway and reduce fertiliser costs. Keywords: Catfish, fishpond waste, pollution, nutrients. Introduction Waste from intensive catfish (Pangasianodon hypophthalmus) aquaculture production has become a pollutant of surface waters in the Mekong Delta, Vietnam (Phuong, 1998). From these ponds, large quantities of liquid and solid waste are discharged to waterways without treatment. Consequently, the pollution of canals or rivers by loading of fishpond waste, rich in nutrients (especially nitrogen, phosphorus and potassium) has emerged as a major concern. Catfish culture in the Mekong Delta has been practiced for a long time but this industry became important for export only after the year 2000 with an annual growth rate of about 15-20 %. Total catfish production in the Mekong delta has increased sixfold from 400,000 tonnes in 2004 to over 1.5 million tonnes in 2007 from ponds that cover about 5,000 ha in the Mekong delta, Vietnam (Phuoung et al. 2008). From the production of these large quantities of fish, it is estimated that about 450 million cubic metres of solid and liquid waste from fishponds is discharged annually directly to water sources (Phuong, 1998). Pollution due to fishpond waste is attributed to high organic carbon and nutrients (Pillay, 1992). The quantity of waste produced depends upon the quantity and quality of feed (Cowey and Cho, 1991). However, integration of aquaculture into existing agricultural systems has been reported to improve productivity and ecological sustainability through better management and improved soil fertility arising from waste recycling (Bartone and Arlosoroff; 1987). Moreover, properly managed composts can reduce the need for fertilisers (Falahi-Ardakani et al. 1987). The nutrients supplied in fishpond solid waste need to be carefully managed in rice fields to avoid significant change in the soil loading of available nutrients. The accumulation of P in soils may over time lead to eutrophication of surrounding waterways, as has occurred in many parts of the world (Brookes et al. 1997). Moreover, excessive N supply to rice crops from the combination of N in solid waste in fertiliser supply may lead to lodging of rice that decreases harvestable grain yield. Hence any scheme to use fishpond solid waste needs to carefully account for the extra nutrients supplied and make appropriate adjustments to fertiliser rates and time of application. The availability of nutrients in fishpond solid waste also needs to be determined. The present study aims at recycling solid wastes from fishponds by using them in rice cultivation to recover the nutrients and make use of the organic content in wastes. The objective of the study was to determine the fertiliser substitution value of the solid waste in order to determine how to adjust recommended fertiliser rates for rice. Materials and methods Solid waste from fishponds in the form of sludge, with up to 60 % water content, was drained and then incubated to allow partial composting. The composition of solid waste for the wet (Cw) and dry season (Cd) is shown in Table 1. Inorganic fertilisers used for field experiments were urea, superphosphate and muriate of potassium. Field experiments on recycling of solid waste were carried out on six consecutive rice crops commencing with the wet season 2007 and ending with the dry season 2010 at the Cuu Long Rice Research Institute farm at O Mon, Can Tho Province (soil type Umbri-EndoOrthiThionic-Gleysols). Soil characterisation is given in Table 2. Treatments comprised inorganic fertiliser (T1-control) at the recommended dosage of 60N-17.44P- 49.8K/ha for wet season and 80N-17.4P-49.8K/ha for dry season crops, respectively. Fishpond solid waste was applied at 1, 2 or 3 tonnes/ha on dry weight basis in combination with inorganic fertiliser dosages of 1/3 (referred to as treatments T2, T3, T4) or 2/3 (referred to as treatments T5, T6 and T7, respectively) of those applied in the control. Experiment was laid out in randomized block design with three replications and plot size of 7x7 m. Direct seeding of short duration rice cv. Thai Bonet was used for both wet and dry season crops. All fishpond solid waste was applied before planting as was 50 % of the inorganic P and K. The remaining P and K was applied at panicle initiation stage at 35 days after sowing (DAS) while N was split 3 times (7, 20 and 35 DAS) with 25, 50 and 25 % applied, respectively. Water level was maintained at 2 cm depth throughout the crop cycle. Yield components were measured on samples collected in two quadrats of 0.5x 0.5 m. Actual yields were recorded by harvesting 5 m 2 in every plot. Rough rice was then dried, weighed and measured for moisture content. Manual harvesting involved cutting the upper 2/3 of rice plant from the base as is conventional practice by farmers. Threshing was carried in the rice fields leaving rice straw in situ. Under triple rice pattern, straw is usually spread evenly and then burned to facilitate land preparation by rotary tillering for the next crop. However, there is still 1/3 of rice straw left on paddy under double rice system because timing is not so strict and ploughing can be carried out when rice stalks are present on the paddy. Organic carbon is determined by wet digestion; analysis of nutrients (N, P, K, Ca, Mg, Fe, Cu, Zn, Mn) followed standard methods for soil (Page et al. 1982), plant analysis (Chapman and Pratt, 1961); water and wastes samples analysis followed methods for chemical analysis of water and wastes (MCAWW) EPA/600/4/79-020 revised March 1983. Statistical analysis was completed with IRRISTAT software version 5.1 by applying a balanced one-way ANOVA. Nutrient (N, P, K) balances were calculated following the approach of Dobermann and Fairhurst (2000) to estimate total input and output. Values from Dobermann and Fairhurst (2000) were replaced where possible with locally relevant values. Nutrient budgets for nitrogen, phosphorus and potassium under the double rice system were calculated for the scenario where 2/3 of the straw is removed, which is current practice, and for 100 % retention of straw as an indication of the consequences of different straw management strategies. Results In the wet season 2007, rice yields were not significantly different among the treatments. However, due to the uniformly low yield ranging from 2.04 to 2.40 t/ha nutrients in this season were probably not limiting factors. Rice yields increased to 6 t/ha in the dry season 2008 (Fig. 1). Treatment T1 (100 % inorganic fertiliser at recommended rate for dry season) achieved the highest yield. However, it was not significantly higher than treatments T2, T5, T6 and T7. The lower yield in T3 indicated that 1 t of sludge/ha and a reduction in fertiliser by 1/3 resulted in inadequate nutrients for optimal yield. However, an increase in solid waste application rate to 2 or 3 t/ha offset the effects of 1/3 reduction in fertiliser. Moreover, the 2/3 reduction of fertiliser with 1 t of solid waste had not significant effects on yield. Analysis of soil, straw and grain for concentration of macro, secondary and micronutrients showed no variation among treatments for both crops (only macro nutrients analysis were shown in Tables 4-9). This indicated that the use of fishpond solid waste for rice cultivation did not negatively affect rice growth. The highest rice yield was recorded in treatment T7 during wet season 2008 (crop 3) but it was not significantly different from other treatments. There were also no differences in nutrients concentrations in soil, straw and grain analysis. The following dry season crop (4 th ) also had no differences in yield and nutrients concentration among treatments. Nevertheless total nitrogen and available phosphorus in soil were high in treatment T7 and T1, respectively. The highest rice yield in treatment T6 was recorded in the wet season 2009 and it was significant different from others. Meanwhile the lowest yield was found in treatment T2 receiving the lowest fertilization but it was not significantly different to treatment T4. Again treatments T1, T3, T4, T5 and T7 were not statistically different in rice yields. Nitrogen concentration in straw of T6 was also the highest; however, it was not significant different from treatments T1, T3, T5, T7. Potassium concentration in straw of T4 was the lowest in comparison with other treatments. In contrast, T1 had the highest K concentration but it was not significant different with treatment T2, T6 and T7. Again the K concentrations of T6&T7 were more or less the same as T3&T5. In the dry season 2009-2010 (6 th crop), there were no differences in rice yields amongst different treatments even though T7 was the highest. Nitrogen concentration in straw of T2 was the lowest. This data again suggested that low fertilization under this treatment could not meet crop demands for rice growth and development. Nutrient budgets Nitrogen balances over six succeeding crops were presented in Table 11a&b commencing with crop 1 in the wet season 2007 and ending with crop 6 of the dry season 2009-2010. Data in these tables indicated that treatments receiving high N fertilizer (T1, T3, T5, T7) had positive N balances even when straw was removed. When rice straw was returned to paddy completely, treatment T6 also had positive balance in N due to low nutrient requirements of the wet season rice crop. In addition, high N supply with both inorganic and organic forms caused positive N balances in all treatments for the other two wet season crops in 2008 and 2009 even when rice straw was removed. Overall, results indicate that the higher the N input, the higher the positive N balance. Rice yields in dry season crops were about 2 times higher than wet season crops indicating that nutrient removal will be about 2 times higher; consequently, N balances for this crop under straw removal were mostly negative except for treatments T5 and T7 of crop 6 because they were received high dosages of manure and N fertilizer. In the cases where rice straw was fully retained, there were outstanding positive N balances of treatments T1, T3, T5, T7 and also T6 in the 6 th crop. Balances in phosphorus over 6 continuous rice crops were always positive even in the case of straw removal. This indicated that fertilisers and solid waste dosages of this experiment were higher than crop removal. Phosphorus might build up in this acid soil over long time use with both the present P fertiliser application and if solid waste was applied regularly (Table 12 a&b). When straw was removed, K balances in wet seasons were mostly positive except in T2&T4 in the first two crops due to low K application. This trend was reversed in dry season rice crops due to high yields as a consequence of high nutrient requirements. Since treatments T1 and T7 at crop 4 th had received high K dosage either in inorganic or organic forms, they were still positive in K balances. When rice straw was returned to paddy, K balances over all treatments were positive. This confirmed that rational use of rice straw either by retention in paddy fields or by making compost or mixing with fishpond solid waste can help farmers save money for K fertilisers. Changes in soil properties The most impressive change in chemical properties was the organic carbon content in soil of treatment T7 that had increased after crop 2 nd (Table 14). From there on carbon content in soil under this treatment did not increase further. Total N and K were also increased substantially over time, with the use of fertiliser and fishpond waste after 6 subsequent crops. Zinc content in soil increased significantly resulting from high Zn content in fishpond waste application to paddy. Discussion Rice production in the Mekong delta is mainly monoculture rice under double or triple cropping per year. Wet season rice has lower yield than dry season crops (Hoa 2006). Recent study indicated that organic carbon accumulated in paddy under continuous submergence but anaerobic decomposition of debris will also inhibit N mineralization (Olk et al. 2000). Ve et al. (1993) showed that triple rice might have higher total N in soils than double rice but N mineralization was very low. Results in this study also indicated that total N was increased. Negative N balance mainly occurred in dry season crops (T2&T4) in treatments having low N supply indicating that these combinations were not sufficient to maintain sustainable rice production even in the case where rice straw was fully returned to the paddy fields. Nitrogen balances in these studies also pointed out that N fertiliser in the wet season can be reduced further on account of low yield potential to alleviate pollution risk. Alternatively limiting factors must be identified to increase rice yield in the wet season in order to use fertilisers more efficiently. Survey data by Tan et al. (2000) revealed that most of farmers in the Mekong delta applied incorrect fertiliser dosages for wet season crops. They normally used about 123 kg N/ha for wet season rice crops but only 113 kg N/ha for the dry season even though yield in the wet season was lower. The reason behind this choice was that rice in the wet season is stunted and farmers only know the application of nitrogen as a method to increase rice plant health. Hence the risk of positive N balances in farmers’ rice fields may be greater than that calculated here on account of greater wet season N fertiliser application by farmers. Long term effects of cropping systems on N balance are still limited and giving contradictory results. Campbell and Zentner (1993) found negative N balances after 24 years of crop rotation but Drinkwater et al., (1998) discovered positive N balance on legume-based cropping. Anh (2001) concluded that there were negative N balances in most of soils in Vietnam but he did not give more details to justify these conclusions. These finding may only be true in the case of low fertilization rates, high yielding crops and complete removal of crop residue. Data in Table 11a&b consolidated this explanation. Pampolino (2007a) reported that total N in soil changed very little or not at all after 13 years under rice cultivation without fertilization. He pointed out that N loss was far higher than N fixation when N fertiliser was applied at high dosage. An experiment at CLRRI on ammonia volatilization with 100 kg N/ha were set up in 2009 on a paddy field. Results gave out NH 3 loss at only 1 kg N/ha for the wet season and 11 kg N/ha in dry season rice crops (Giau, 2010). These figures were used to adjust N balance of the present study but the change in N balance would not be great. Based on data of N balances over all 6 crops under different treatments in this study, it might be concluded that the treatment T1 (recommended dosage of inorganic fertilisers) used in this study was reasonable to maintain N balance when straw was removed. The treatment combination of T3 or T6 could be recommended to farmers who could prepare manures for their own use to save money on fertiliser costs. Further reduction in inorganic fertilisers might be possible when all straw was retained and in this case treatments T2 &T4 are recommended. Phosphorus balances (Table 12a&b) showed that only treatments T2, T4 and T6 (low inorganic fertilization) in the first dry season crop (crop 2 nd ) had negative P balances. The other 5 rice crops had positive P balances. This finding was similar to the results of Giau (2010) studying P balances for the rice-rice system on Mekong delta soils. Dat (2009) also found positive P balances on the rice-maize-rice system. Over 2 wet season rice crops, the 5 th crop compared to 3 rd crop, the available P over all treatments was significantly increased (Table 15). Treatments T2, T6 and T7 after the 5 th crop were statistically higher than those by the end of the 3 rd crop (Table 15). These results suggest that soil amended with fishpond solid waste could increase available P on this acid soil. Since the present available P levels are still quite low, it will take some time before there is sufficiently high P levels to replace the need for fertiliser application or to create a risk of off-site effects of P from the continual use of fishpond waste. However, as a precaution, and to minimise costs of rice production there appears to be ample scope for substantial decreases in P fertiliser application when fishpond waste is applied. Potassium balances were positive when straw was completely returned to paddy and also for those treatments receiving high K fertilization, even with straw removal (Tables 13 a&b). These findings were similar to Hoa (2006) who studied K balances on a CLRRI soil. Doberman et al. (1998) stated that most intensively cultivated paddy fields in Asia had negative K balance. Potassium balance depended on many factors such as water source, K adsorption by soil, straw management and rice yields. Another investigation on double rice farming in the Mekong delta also showed positive K balance for exchangeable, non-exchangeable and total K in soil (Giau, 2010). Overall results indicated that farmers in the Mekong delta should make greater use of rice straw and fishpond solid waste to return K to their paddy for sustainable rice cultivation and to reduce costs for rice production. [...]... Toulouse, France Phuong, N.T., Oanh, N.T.H., Tuan, N .A. , 2008 Striped Catfish (Pangasianodon hypophthalmus) Aquaculture in Vietnam: An Unprecedented Development within a Decade Catfish Aquaculture in Asia: Present Status and Challenges for Sustainable Development Handbook and Abstracts from Conference at CanTho University, CanTho City, Vietnam p 25 Pillay, T.V.R 1992 Aquaculture and Environment Blackwell... Sat, C.D, Castillo, E.G., Singh, U., 1995 Effect of phosphorus and growing season on rice growth and nutrient accumulation on acid sulfate soils, in: Vietnam and IRRI: A Partnership in Rice Research International Rice Research Institute, Manila 1099, Philippines pp 123-135 Cripps, S.J 1995 Serial particle size fractionation and characterisation of an aquacultural effluent Aquaculture 133, 323-339 Falahi-Ardakani,... rice paddy area Greater than 60 ha per ha of fishpond area would be advisable to minimise the risks of nutrient build up as discussed above and to allow for the unavailability of some fields at the time when the solid waste was available Since about 5,000 ha of land is occupied by fishponds in the Mekong delta, > 300,000 ha of padi land in close proximity to the fishponds may be required to treat solid. .. environmental water quality Acknowledgements This research was financially supported by CARD project VIE/023/06 The assistance of staff in the Soil Science Department and a student of An Giang University to carry out this study are greatly appreciated Thanks also to Cuu Long Rice Research Institute and the Ministry of Agriculture & Rural Development, Vietnam for the facilities and services granted to... Chapman, H.D., Pratt, P F., 1961 Methods of analysis for soil, plant and water Division of Agricultural Sciences, University of California, Riverside Cho, C.Y., Hynes, J.D., Wood, K.R., Yoshida, H.K., 1991 Quantification of fish culture wastes by biological and chemical (limnological) methods, in: Cowey C.B and Cho C.Y (Eds), Nutritional Strategies and Aquaculture Waste University of Guelph, Canada...Data in this studies had revealed that organic carbon as well as total N built up after 6 crops continuously amended with fishpond solid waste (Table 14) This will benefit soils with very low organic carbon content especially in areas of the closed dike system of An Giang province under triple rice cropping sequence where current total fertiliser application /crop is about 600-700 kg/ha Solid waste... significant concern except before direct sowing of rice seeds on the prepared seedbed Assuming a fish harvest of 300 t/ha/yr from fishponds, and a feed conversion of 1 tonne of fish biomass for every 1.6 t of feed, 1 ha of fishpond generates about 180 t of organic waste Based on an application rate of 3 t/ha, about 60 ha of padi land per 1 ha of fishpond This represents a minimum ratio of fishpond area to... Straw 13.5 1.8 31.4 HI 0.5 from Dobermann and Fairhurst (2000) OUT3 Percolation 17 1 10 Dobermann and Fairhurst (2000) Gaseous OUT4 losses 1 0 0 Gaseous loss by NH3 volatilization and denitrification 86.4 10.8 48.9 17.6 11.5 26.9 Straw removed (only 2/3) 31.1 13.2 58.2 Straw retained 100% Net balance Table 1 1a: Balance for N in each crop with full, 1/3 and 2/3 fertiliser rates applied (Straw removal)... (Ipomoea aquatica) with these two treatments were not statistically different The application of fishpond solids can cause “clogging” of soil pores at the soil surface, due to the organic and inorganic particles applied Clogging interferes with the movement of gases and liquids into the soil matrix (Fuller and Warrick 1985; Loehr et al 1979) For rice, exact levelling is required to prevent waste accumulating... (control) –inorganic fertiliser at the recommended dosage of 60N-17.44P-49.8K/ha for wet season and 80N-17.4P-49.8K/ha for dry season crops, respectively Fishpond sludge compost was applied at 1, 2 or 3 tonnes/ha on dry weight basis in combination with inorganic fertiliser dosages of 1/3 (referred to as treatments T2, T4, T6) or 2/3 (referred to as treatments T3, T5 and T7, respectively) of those applied in . cv. Thai Bonet was used for both wet and dry season crops. All fishpond solid waste was applied before planting as was 50 % of the inorganic P and K. The remaining P and K was applied at panicle. Final Nutrient recovery by rice crops as a treatment for aquaculture solid waste: crop yield, nutrient status and nutrient budgets Cao van Phung 1 1. Cuu Long Rice Research Institute,. Ca, Mg, Fe, Cu, Zn, Mn) followed standard methods for soil (Page et al. 1982), plant analysis (Chapman and Pratt, 1961); water and wastes samples analysis followed methods for chemical analysis